key: cord-0821033-xcbaccc7
authors: Williams, John; Petrik, Leslie; Wichmann, Janine
title: PM(2.5) chemical composition and geographical origin of air masses in Cape Town, South Africa
date: 2020-10-07
journal: Air Qual Atmos Health
DOI: 10.1007/s11869-020-00947-y
sha: 40b7fb5acf764bd7102af9496f2d95c6fad39b4d
doc_id: 821033
cord_uid: xcbaccc7

PM(2.5) in the indoor and outdoor environment has been linked in epidemiology studies to the symptoms, hospital admissions and development of numerous health outcomes including death. The study was conducted during April 2017 and April 2018. PM(2.5) samples were collected over 24 h and every third day. The mean PM(2.5) level was 13.4 μg m(−3) (range: 1.17–39.1 μg m(−3)). PM(2.5) levels exceeded the daily World Health Organization air quality guideline (25 μg m(−3)) on 14 occasions. The mean soot level was 1.38 m(−1) × 10(−5) (range: 0 to 5.38 m(−1) × 10(−5)). Cl(−), NO(3)(−), SO(4)(2−), Al, Ca, Fe, Mg, Na and Zn were detected in the PM(2.5) samples. The geographical origin of air masses that passed Cape Town was estimated using the Hybrid Single Particle Lagrangian Integrated Trajectory software. Four air masses were identified in the cluster analysis: Atlantic-Ocean-WSW, Atlantic-Ocean-SW, Atlantic-Ocean-SSW and Indian-Ocean. The population of Cape Town may experience various health outcomes from the outdoor exposure to PM(2.5) and the chemical composition of PM(2.5). ELECTRONIC SUPPLEMENTARY MATERIAL: The online version of this article (10.1007/s11869-020-00947-y) contains supplementary material, which is available to authorized users.

Various indoor and outdoor air pollutants are linked in epidemiology studies to the symptoms, hospital admissions and development of numerous health outcomes such as asthma (Fan et al. 2016) , cardiovascular disease (Cesaroni et al. 2014; Wang et al. 2015; Münzel et al. 2018) , skin diseases (Balmes 2019) , birth outcomes (Li et al. 2019 ), sperm quality (Lafuente et al. 2016) , type 1 and 2 diabetes (Ritz et al. 2019; Howard 2019) , lung cancer (Lipfert and Wyzga 2019, Hamra et al. 2014 )-even with the spread and increase of Covid-19's morbidity and mortality (Bilal et al. 2020; Comunian et al. 2020 ; Rodríguez-Urrego and Rodríguez-Urrego 2020) and other disease mortality (Fajersztajn et al. 2017; Liu et al. 2019; Orellano et al. 2020 ). Most of these epidemiology studies were conducted in the developed world and very few in Africa (Ostro et al. 2018 ; Rodríguez-Urrego and Rodríguez-Urrego 2020, Orellano et al. 2020; Liu et al. 2019; Ofori et al. 2020 , Katoto et al. 2019 Wichmann and Voyi 2012; Coker and Kizito 2018; Lokotola et al. 2020 ).

An epidemiology study in Cape Town, South Africa, reported that exposure to outdoor particulate matter smaller or equal to 10 μm in aerodynamic diameter (PM 10 ), nitrogen dioxide (NO 2 ), sulphur dioxide (SO 2 ) levels in Cape Town during 2001-2006 posed a much higher risk to die from cardiovascular and respiratory diseases than reported in developed countries, even though the outdoor levels were on average similar to those in European cities (Wichmann and Voyi 2012) .

Another study in Cape Town observed that a 10 μg m −3 increase in PM 10 , NO 2 , SO 2 led to increases in 2.4% (1.3%, 3.5%), 5.1% (3.0%, 7.2%) and 5.1% (3.0%, 7. 2%) in cardiovascular disease hospital admissions during 2011-2016, respectively (Lokotola et al. 2020) . These adverse effects were stronger on days warmer than 20.3°C. Wichmann and Voyi (2012) and Lokotola et al. (2020) did not investigate particulate matter smaller or equal to 2.5 μm in aerodynamic diameter (PM 2.5 ) as this air pollutant is not currently monitored in Cape Town. The daily and yearly PM 2.5 South African national ambient air quality standard came into effect on June 29, 2012 (Department of Environmental Affairs Electronic supplementary material The online version of this article (https://doi.org/10.1007/s11869-020-00947-y) contains supplementary material, which is available to authorized users. 2012). It is widely accepted that PM 2.5 is more hazardous to human health than PM 10 , as it can penetrate deeper into the respiratory tract than PM 10 , penetrate the lung barrier and enter the blood system (World Health Organization 2013) .

Very few studies in Africa reported on PM 2.5 levels (Maenhaut et al. 1996; Petkova et al. 2013; Gaita et al. 2014; Snider et al. 2016; Fayiga et al. 2018; Tshehla and Djolov 2018; Kalisa et al. 2019; deSouza 2020) . No study ever reported on PM 2.5 levels in Cape Town nor investigated its seasonal and weekly variation, chemical composition and possible source region contributions by using backward trajectory cluster analysis. The objectives of this study were to address these research gaps.

The sampling site was at an urban background, located on the roof of a house in the suburb of Kraaifontein, Cape Town (3 m above ground level, 27 km ENE of the city centre and 1 km from a busy freeway) ( Fig. 1 and Fig. S1 ). This site was a favourable choice for sampling due to the assurance of safety and a continuous supply of electricity. The University of the Western Cape campus was not selected as sampling site due to its close proximity to Cape Town International Airport.

Cape Town occupies the south-western most point of the Western Cape Province. Topographically, the city is situated 10-150 m above sea level and has many peaks exceeding 300 m, the most well-known being Table Mountain (1000-1100 m above sea level) .

Cape Town has a Mediterranean-style climate that is influenced by both the warm Agulhas current and the cold Benguela current (Western Cape Air Quality Management Plan 2016; Beck et al. 2018; World Meteorological Organization 2020) . It is the second-most populous city in South Africa; 3.7 million residents during the latest census of 2011 (Western Cape Air Quality Management Plan 2016). PM 2.5 sampling, gravimetric and chemical analyses 24-h ambient PM 2.5 filter samples were collected manually every third day for a period of 1 year (April 18, 2017 , to April 16, 2018 using GilAir-5 personal air samplers (Sensidyne, Schauenburg Electronic Technologies Group, Mulheim-Ruhr, Germany) on 37 mm PTFE membrane filters (Zefon International, Florida, USA). The flow rate was 4 l/min, similar to other studies (Gaita et al. 2014; Novela et al. 2019; Adeyemi 2020) . Sampling started 9 a.m. and ended 9 a.m. the next day. The start and stop times were selected for practical reasons as starting and stopping a sample at midnight was not practical. PM 2.5 was sampled on the same days and times in Pretoria and Thohoyandou, South Africa (Novela 2019; Adeyemi 2020) . A large multi-country study started and ended sampling at 9 a.m. to reduce loss of semi-volatile components (Snider et al. 2016) . Snider et al. (2016) described that the loss rates of NH 4 NO 3 during passive air flow were less than during active air flow. The sampling protocol of Snider et al. (2016) was designed to actively sample for one diurnal cycle and to avoid daytime sampling after collecting night time PM 2.5 .

Other studies used pumps that were similar to the GilAir-5 for ambient air monitoring (Novela 2019; Adeyemi 2020; Mwase 2020). Mwase (2020) indicated that there was a good correlation between PM 2.5 levels measured on filter samples using a GilAir-5 pump and those obtained using a continuous real-time instrument in Pretoria, South Africa during May 2018 to May 2019 (Fig. S2 ).

In total, 146 24-h PM 2.5 filter samples (including 25 duplicate samples) were collected on 121 days during the 1-year study period. In addition to the 24-h PM 2.5 filter samples, four composite samples (two weekdays and two weekend days) were collected over four consecutive weeks (9 am to 9 am at intervals of 7 days) during September 2017 and January 2018 to determine the anion and elemental composition of PM 2.5 . Total exposure time for each composite sample was 96 h.

The 24-h PM 2.5 filter samples were weighed at the School of Health Systems and Public Health (SHSPH), University of Pretoria (UP) in batches of 20 before and after sampling. An ultra-micro-balance (Mettler-Toledo XP6) was used under climate-controlled conditions (temperature: 20.1-22.0°C, relative humidity: 43-54%) (Fig. S3 ). These batches were hand delivered and kept dry from direct sunlight and at room temperature during transit.

The 96-h PM 2.5 filter samples were weighed at the Department of Chemical Sciences, University of the Western Cape (UWC) with a microbalance (Mettler-Toledo ML 204) before and after sampling.

The 24-h and 96-h PM 2.5 filter samples were stored in a refrigerator at 4°C. After gravimetric analysis, reflectance measurements were performed using an EEL43 reflectometer (Diffusion Systems Ltd. EEL model 43 D) at the SHSPH, UP. Measuring light absorption or reflectance of PM collected on filters is an alternative method to determine elemental carbon, a marker for particles produced by incomplete combustion; also referred to as soot (RUPIOH 2002) .

The results were transformed into absorption coefficient (hereafter 'soot'). The following equation was used, as done in other studies (RUPIOH 2002; Cesaroni et al. 2014 ):

where a is the absorption coefficient (m −1 × 10 −5 ), V the sampled volume (m 3 ), R 0 the reflection of a primary control filter (%), R f the reflection sampled filter (%) and A the loaded filter area (m 2 ). The average reflectance of the primary control filter was 100.075 (SD 0.1). Soot levels (m −1 × 10 −5 ) of the 96-h PM 2.5 filter samples were converted to equivalent black carbon (eBC) levels (μg m −3 ) in order to calculate the percentage mass in comparison with PM 2.5 mass. The following equation was used, as done in other studies (Davy et al. 2017) :

where A is the loaded filter area (8.55 × 10 −4 m 2 ), V the sampled volume (m 3 ), σ ATN is black carbon extinction coefficient (19.5 m 2 g −1 for PTFE filters), k is the loading correction factor (0.3 for PTFE filters) and R is reflectance. Elemental levels of the 96-h PM 2.5 samples were determined at UWC using a Varian 710-ES Inductively Coupled Plasma-Optical Emission Spectrometer (Supplementary text S1). Al, Ca, Fe, Mg, Na and Zn levels were above the LOD (0.001 μg m −3 ), whilst As, Be, Cd, Cr, Co, Cu, Pb and Li levels were below the LOD.

Anion levels of the 96-h PM 2.5 filter samples were determined using a Dionex ICS-1600 Ion Chromatograph at UWC 

The geographical origin of air masses that passed Cape Town was applied as surrogates for long-range transported air pollution from distant sources and its composition, as done in other studies (Kim et al. 2014; Saikat et al. 2015; Schwarz et al. 2016; Molnár et al. 2017; Tshehla and Djolov 2018; Novela 2019; Adeyemi 2020) .

For each day in the 1-year study period, 72-h backward trajectories were produced using the Hybrid Single Particle Lagrangian Integrated Trajectory software (HYSPLIT) (the latest version, July 2018, was downloaded at www.ready. noaa.gov/HYSPLIT.php).

The HYSPLIT software downloaded and executed by the NCEP/NCAR (National Centers for Environmental Prediction/National Centre for Atmospheric Research) Global Reanalysis Meteorological Data at the web server of the National Oceanic and Atmospheric Administration Air Resources Laboratory (NOAA ARL). An analysis field (resolution 2.5°× 2.5°and 17 vertical levels) was provided every 6 h (0:00, 6:00, 12:00, 18:00) for a 72-h backward trajectory and the wind field was interpolated linearly between each analysis, as done in other studies (Wichmann et al. 2014; Molnár et al. 2017 ; Novela 2019; Adeyemi 2020).

Since a single backward trajectory has a large uncertainty and is of limited significance, an ensemble of trajectories with 500 m starting height and a fixed offset grid factor of 250 m was used in this study (i.e. 250 m and 750 m also used) as done in other studies (Wichmann et al. 2014; Molnár et al. 2017 , Novela 2019 , Adeyemi 2020 .

A total of 4380 72-h backward trajectories were generated and applied in the cluster analysis with the HYSPLIT software. Four geographical origins of air masses were identified in the cluster analysis ( Fig. 2, Fig. S4 and Fig. S5 ): Atlantic-Ocean-WSW, Indian-Ocean, Atlantic-Ocean-SW and Atlantic-Ocean-SSW. Each day in the 1-year study period was allocated to one of these geographical origins of air masses as done in other studies (Wichmann et al. 2014; Molnár et al. 2017 , Novela 2019 , Adeyemi 2020 ).

Additionally, existing air pollution data were obtained from the City of Cape Town after the PM 2.5 sampling campaign had ended. The hourly data included daily levels of PM 10 , NO 2 , SO 2 and ground-level ozone (O 3 ) measured at six ambient air quality monitoring (AAQM) stations during the 1-year study period. The National Environmental Management: Air Quality Act (NEMAQA) (Act 39 of 2004) requires the monitoring of criteria air pollutants in South Africa (Department of Environmental Affairs 2005). The NEMAQA currently enforces NAAQS for PM 2.5 , PM 10 , NO 2 , SO 2 , carbon monoxide, ground-level O 3 , lead and benzene (Department of Environmental Affairs 2005 , 2012 . However, as mentioned before, PM 2.5 is not currently measured at any AAQM station in the City of Cape Town. Figure 1 indicates the location of the six AAQM stations in the city (Supplementary text S3 and S4; Table S7 ). The AAQM stations at Wallacedene, Goodwood, Tableview, City Hall and Somerset-West are within a 30 km radius of the PM 2.5 sampling site in Kraaifontein. The PM 10 , NO 2 , SO 2 , O 3 levels measured at these five AAQM stations were used to indicate potential local sources of ambient PM within a 30 km radius of the PM 2.5 sampling site. The Atlantis AAQM station is situated 37 km from the PM 2.5 sampling site and 100 km from the town of Saldanha, which has ore refineries. The Atlantis AAQM station was used to indicate longrange transported PM 2.5 that arrived at the PM 2.5 sampling site.

These six AAQM stations continuously assess real-time levels of the criteria air pollutants using equivalent methods of the United States Environmental Protection Agency and in accordance with ISO 17025 guidelines (Department of Environmental Affairs 2005; Western Cape Air Quality Management Plan 2016).

Hourly temperature (°C), relative humidity (%), wind speed (m s −1 ) and precipitation (mm) data were obtained from the South African Weather Service for the 1-year study period.

The daily averages of PM 10 , NO 2 , SO 2 , ground-level O 3 and meteorological variables were calculated from 9 a.m. to 9 a.m. on days when PM 2.5 was sampled. The daily averages were based on at least 18 hourly values. If more than six hourly values were missing during the 24-h period, then the daily average was set as missing.

Statistical analyses were performed with SAS version 9.3. Descriptive statistics were reported for the 121 observations According to the Shapiro-Wilk's test, in general, the 121 observations of 24-h air pollution and meteorological variables did not have normal Gaussian distributions and nonparametric tests were applied. Spearman rank-ordered correlation analyses were applied to investigate the correlation between the 24-h air pollution and meteorological variables for the 1-year study period and by seasons.

Seasons were defined as: autumn (18/4/2017 to 31/5/2017 and 1/3/2018 to 16/4/2018), winter (1/6/2017 to 31/8/2017), spring (1/9/2017 to 30/11/2017) and summer (1/12/2017 to 28/2/2018).

Kruskal-Wallis tests were conducted to determine whether the 24-h median air pollution levels differed significantly between seasons and between the four geographical origins of air masses. Wilcoxon's rank-sum test was applied to test whether 24-h median air pollution levels differed significantly between weekdays and weekends.

Descriptive statistics are presented in Table 1 . Time-series graphs of PM 2.5 , soot and the meteorological conditions are presented in Fig. 3 . The mean temperature was 17.7°C and ranged from 9.2 to 25.3°C. Wind speed ranged from 1.0 to 8.1 m s −1 and relative humidity 37.3 to 90.7%. Figure S6 indicates the frequency of wind speed by seasons and direction. There was a severe drought in Cape Town during the sampling period and the maximum precipitation recorded was 11.4 mm (Fig. S7) .

The mean PM 2.5 level for the 1-year study period was 13.3 μg m −3 , which was below the yearly South African National Ambient Air Quality Standard (SA NAAQS) (20 μg m −3 ) (Department of Environmental Affairs 2005), but exceeded the yearly WHO air quality guideline (10 μg m −3 ) (World Health Organization 2005). Median PM 2 . 5 levels in winter (13.2 μg m − 3 ) and spring (18.0 μg m −3 ) were significantly higher (p < 0.05) than in autumn (9.8 μg m −3 ) and summer (8.9 μg m −3 ). The daily WHO air quality guideline (25 μg m −3 ) was exceeded on 5 and 9 days during winter and spring, respectively. The daily SA NAAQS (40 μg m −3 ) was never exceeded. These exceedances indicate that the population of Cape Town may experience various health outcomes due to outdoor PM 2.5 exposure, as indicated previously.

The median PM 2.5 level on 38 weekend/public holidays (14.1 μg m −3 ) was significantly higher (p < 0.05) than that on 83 weekdays (9.9 μg m −3 ). A possible reason may be that neighbours close by performed metal works over weekends or due to the South African tradition of barbequing on weekends; the samples were collected in a residential area. However, No missing values for PM 2.5 or soot. 1 and 7 missing values for relative humidity and wind speed, respectively median soot levels on weekdays and weekends did not differ significantly, see below.

The mean PM 2.5 level in this study was lower than the mean in 499 cities of 24 countries (37.5 μg m −3 ) (Liu et al. The mean soot level was 1.368 m −1 × 10 −5 (Table 1) . Median soot levels in autumn (1.493 m −1 × 10 −5 ) and winter (2.008 m −1 × 10 −5 ) were significantly higher (p < 0.05) compared with those in spring (0.837 m −1 × 10 −5 ) and summer (0.547 m −1 × 10 −5 ). Soot levels had a consistent downward trend during June 2017 to December 2018 (Fig. 3 ). Autumn and winter had the largest variations in soot levels. Median soot levels on weekdays (0.916 m −1 × 10 −5 ) and weekends (1.096 m −1 × 10 −5 ) (p > 0.05) did not differ significantly. There is no SA NAAQS or WHO air quality guidelines for soot.

Very few studies in Africa reported soot levels. The mean soot levels in Pretoria were higher and varied between 2.3 m −1 × 10 −5 during April 2017 to April 2018 and 0.02 m −1 × 10 −5 during May 2018 to Apr 2019 (Adeyemi 2020, Mwase 2020). The mean soot levels in Thohoyandou, a town located in a rural area about 2000 km north of Cape Town, were lower: 0.69 m −1 × 10 − 5 during April 2017 to April 2018 (Novela 2019). Luben et al. (2017) concluded in a review that atmospheric black or elemental carbon is a risk factor for hospital admissions and mortality. Cesaroni et al. (2014) focused on air pollution exposure over many years and reported a 10% increase in acute myocardial infarction or other acute and sub-acute forms of ischemic heart disease per unit m −1 × 10 −5 increase in soot levels in five European countries.

The 96-h PM 2.5 mass ranged between 300 and 400 μg ( Table 2 ). The 96-h PM 2.5 level was higher on Saturdays (17.4 μg m −3 ) than on Thursdays (13.0 μg m −3 ) in September 2017 (spring). In contrast, the 96-h PM 2.5 level was lower on Saturdays (13.0 μg m −3 ) than on Tuesdays (17.4 μg m −3 ) in January 2018 (summer). The meteorological conditions were similar during the 24-h and 96-h sampling.

The largest fraction of PM 2.5 was due to anionic and metallic species ranging from 31 to 54% of mass and 27-51% of mass, respectively (Table 2 and Fig. S8 ). Na and Cl − were the most abundant constituents of PM 2.5 . The Atlantic Ocean (20 km west from the study site) and Indian Ocean (25 km south from the study site) are the most probable sources of Na and Cl − in the PM 2.5 samples. Several epidemiology studies that investigated acute health outcomes, such as hospital admissions, published since 2005 have included a source category for sea salt. Sea salt has not been associated with adverse health outcomes (World Health Organization 2013).

A study from Pretoria, located inland about 600 km from the Indian Ocean, sampled PM 2.5 and reported lower mean 24-h Cl − levels during spring and summer, 19.3 ng m −3 and 16.8 ng m −3 , respectively (Adeyemi 2020). A study from Nairobi, Kenya, located inland about 500 km from the Indian Ocean, sampled PM 2.5 and reported lower mean Cl − (Gaita et al. 2014) .

Mg may also originate from sea spray, although it was only detected in the January 2018 samples. Ca was detected in three of the four samples. Ca content can be attributed to either sea sand, soil or mineral dust due to traffic or wind. The mean 24h Ca levels were much lower in Pretoria, namely 95.4 ng m −3 and 87.8 ng m −3 during spring and summer, respectively. Mean Ca levels (0.31 μg m −3 ) were lower in Nairobi, Kenya (Gaita et al. 2014 ). Tshehla and Djolov (2018) reported PM 2.5 Ca levels in a rural area in Limpopo province, South Africa, that ranged from 0.3 to 9.9 μg m −3 .

Samples collected in Saturdays during spring and summer contained Al (0.4-0.7% of mass) and Fe (7.4-9.4% of mass); these elements were not detected in samples collected on Tuesdays and Thursdays. A possible reason for Fe detected in weekend samples is that two neighbours, approximately 20-50 m from the study site, had performed metal works over weekends.

The mean 24-h Fe levels measured at a background site in Pretoria were lower, namely 0.355 μg m −3 and 0.237 μg m −3 , during spring and summer respectively and 20.9 ng m −3 and 9.9 ng m −3 for Zn (Adeyemi 2020) . A study from Nairobi, Kenya, reported lower mean Fe and Zn levels, namely 0.53 μg m −3 and 0.91 μg m −3 , respectively (Gaita et al. 2014 ). Tshehla and Djolov (2018) reported Fe levels that ranged from 0.1 to 1.4 μg m −3 . A large European cohort epidemiology study reported much lower Fe and Zn levels (Beelen et al. 2015) . Even at such lower Fe and Zn levels, an increase of 3% in natural-cause mortality was observed per 500 ng m −3 increase in Fe or per 20 ng m −3 increase in Zn (Beelen et al. 2015) . The observed Fe and Zn levels, if assumed to be experienced citywide in Cape Town, may thus pose a significant risk to human health.

Zn:Al ratios indicate the relative contribution of local road dust to PM 2.5 levels (Snider et al. 2016) . Al is predominantly from natural sources (Snider et al. 2016) , whilst Zn is mainly from tire wear, but also from solid waste or biomass burning and industrial emissions. Snider et al. (2016) reported Zn:Al ratios that ranged from 0.13 to 3.74 with a mean of 0.73. The mean ratio in this study was 2.17, which is higher than of the Pretoria study site (0.86) reported by Snider et al. (2016) . SO 4 2− and NO 3 − were present in all samples and indicated combustion sources in the area, which may include traffic and biomass fuel burning. SO 4 2− in PM 2.5 leads to a substantial increase in the bioavailable metals and soot (World Health Organization 2013). A review concluded that natural-cause mortality increased by 15% and 17% per 1 μg m −3 increase in SO 4 2− and NO 3 − , respectively (Atkinson et al. 2015) . The observed SO 4 2− and NO 3 − levels, if assumed to be representative of levels in Cape Town, may thus pose a significant risk to human health. The inorganic carbon fraction ranged from 7.0-14.2% of mass and the level was higher on Saturdays than on Tuesdays and Thursdays, which may be due to the South African tradition of barbequing on weekends.

Another sizeable part of PM 2.5 mass was the 'undetermined' portion that consisted most probably of ammonium (as NH 4 Cl), volatile organic carbons, polyaromatic hydrocarbons, peroxyacyl nitrates and water (Kreidenweis et al. 2008 ; Widziewicz-Rzońca and Tytła 2020).

Four geographical origins of air masses were identified: Atlantic-Ocean-SW, Atlantic-Ocean-SSW, Atlantic-Ocean-WSW and Indian-Ocean (Fig. 2) . Air masses emanating from the Atlantic Ocean dominated in winter (87%), summer (73%), spring (77%) and the entire year (71%) ( Table S7 ). In autumn, 51% of the air masses emanated from the Indian Ocean, with 29% in the entire study period.

The median 24-h PM 2.5 and soot levels did not differ significantly by the geographical origin of air masses (p > 0.05) ( Table 3) .

The median temperature and relative humidity levels differed significantly by the geographical origin of air masses (p < 0.05) (Table S8) , with the highest temperature (19.7°C) observed when the air mass originated in the warm Indian Ocean and the lowest relative humidity (58.8%) observed when the air mass originated in the cold Atlantic Ocean (Atl-Ocean-SSW). Wind speed and precipitation levels were not influenced by the geographical origin of air masses (p > 0.05).

The correlation between PM 2.5 and soot levels was positive (0.596) (Fig. S9 ) and the strongest during winter (0.818), followed by autumn (0.750), spring (0.546) and summer (0.427) ( Table S9 ). All these correlations were significant.

PM 10 , NO 2 , SO 2 and O 3 levels varied by the hour of the day and indicated possible sources (Figs. S10 to S13; Supplementary text S4). The descriptive statistics are indicated in Table S10 and discussed in Supplementary text S4. ND not detected PM 2.5 and soot levels measured at the Kraaifontein sampling site had positive and significant correlations (p < 0.0001) with PM 10 levels measured 3 km away at the Wallacedene AAQM station (Table 4 ). This may indicate that the PM 10 sources indicated by the Wallacedene AAQM station (Supplementary text S4), namely traffic and biomass burning for space heating and barbequing, may influence the PM 2.5 levels measured at the Kraaifontein sampling site. The correlation between PM 2.5 and PM 10 (0.481) was weaker than the correlation observed in 652 cities in 24 countries (0.78) (Liu et al. 2019) .

PM 2.5 levels had positive and significant correlations with NO 2 levels measured at the Wallacedene, Goodwood, Tableview (18 km away) and City Hall (27 km away) AAQM stations, with the strongest correlations (0.638) between NO 2 levels measured at the Wallacedene AAQM station (Table 4) . NO 2 is a precursor for ions of water-soluble inorganic salts that can partition to the particulate-phase; hence, traffic in the vicinity of these four AAQM stations (Supplementary text S4) may contribute to the PM 2.5 levels measured at the Kraaifontein sampling site. The strength of the correlations with Goodwood, Tableview and City Hall AAQM stations did not follow a clear trend according to distance from the Kraaifontein sampling site. Liu et al. (2019) reported a correlation of 0.48 between PM 2.5 and NO 2 in 652 cities in 24 countries.

As with PM 2.5 , soot levels had positive and mostly significant correlations with NO 2 levels with the strongest correlation (0.726) between NO 2 levels measured at the Tableview AAQM station (Table 4 ). As with PM 2.5 , the strength of the correlations with Goodwood, Tableview and City Hall AAQM stations did not follow a clear trend according to distance from the Kraaifontein sampling site. PM 2.5 levels had positive and mostly significant correlations with SO 2 levels measured at the six AAQM stations, with the strongest correlation (0.597) at the Goodwood AAQM station and the weakest (0.198) at the Atlantis AAQM station (37 km away) ( Table 4 ). As with NO 2 , SO 2 is a precursor for ions of water-soluble inorganic salts that can partition to the particulate-phase; hence, the SO 2 sources indicated by these six AAQM stations (Supplementary text S4), namely traffic and an oil refinery, may lead to higher PM 2.5 levels measured at the Kraaifontein sampling site. The lack of Table S10 significant polluters to the north of the study site and poor correlation with SO 2 levels in the town of Atlantis indicated that air mass transport of airborne particulate matter from the north was minimal. The strength of the correlations did not follow a clear trend according to distance from the Kraaifontein sampling site. Liu et al. (2019) reported a correlation of 0.40 between PM 2.5 and SO 2 in 652 cities in 24 countries. As with PM 2.5 , soot levels had positive correlations with SO 2 levels measured at the six AAQM stations. The strongest correlation (0.681) was between SO 2 levels measured at the Goodwood AAQM station and the weakest (0.231) at the Somerset West AAQM station ( Table 4 ). As with PM 2.5 , the strength of the correlations did not follow a clear trend according to distance from the Kraaifontein sampling site. PM 2.5 and soot levels had negative and mostly insignificant correlations with ground-level O 3 levels measured at Wallacedene and the Goodwood AAQM stations, but a positive and significant correlation with ground-level O 3 levels measured at the Atlantis AAQM station (Table 4) Meteorological conditions can diffuse, dilute and accumulate air pollution. The results are presented in Tables S9 and S11 and discussed in Supplementary text S5.

The mean PM 2.5 level for the 1-year study period was 13.3 μg m −3 , which exceeded the yearly WHO air quality guideline (10 μg m −3 ). Median PM 2.5 levels in winter and spring were significantly higher than in autumn and summer These exceedances indicate that the population of Cape Town may experience various health outcomes due to outdoor PM 2.5 exposure.

Median soot levels in autumn and winter were significantly higher compared with those in spring and summer. The largest fraction of PM 2.5 was due to anionic and metallic species. The inorganic carbon fraction ranged from 7.0-14.2% of mass. Another sizeable part of PM 2.5 mass was the "undetermined" portion.

Four geographical origins of air masses were identified and those emanating from the Atlantic Ocean dominated most of the year. In autumn, the air masses emanated from the Indian Ocean were more prevalent. The PM 2.5 and soot levels did not differ significantly by the geographical origin of air masses though.

It was observed that air pollution sources indicated by the AAQM stations, namely traffic, biomass burning for space heating and barbequing and an oil refinery, may lead to higher PM 2.5 levels measured at the Kraaifontein sampling site.

Recommendations are that all the PM 2.5 samples are analysed for chemical composition to perform source apportionment and health risk assessment studies.

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Acknowledgments The authors express gratitude towards the South African National Research Foundation for funding, the City of Cape Town: Air Quality Division for providing air pollution data, the South African Weather Services for providing meteorological data, Thizwilondi Madzaga and Ilse Wells for assisting with laboratory analyses and Peter Molnár, University of Gothenburg, Sweden, for preliminary feedback during the MSc studies of John Williams.Authors' contributions All authors contributed to the study conception and design. Material preparation, data collection and analysis were performed by all the authors. The first draft of the manuscript was written by John Williams and all authors commented on previous versions of the manuscript.Funding This study is funded by the South African National Research Foundation (Grant CPT160424162937, Janine Wichmann was the PI).Data availability Upon request, but then, the authors want to be coauthors on the other study's manuscript.

Conflict of interest The authors declare that they have no conflict of interest.